SORPTION KINETICS OF Pb (II) AND Cd (II) IONS VIA BIOMASS SURFACE OF PLANTAIN PEEL WASTE

www.arpapress.com/volumes/vol13issue2/ijrras_13_2_29.pdf SORPTION KINETICS OF Pb (II) AND Cd (II) IONS VIA BIOMASS SURFACE OF PLANTAIN PEEL WASTE A.K. Asiagwu Department Of Chemistry, Delta State University, Abraka, Nigeria drasiagwu@yahoo.com ABSTRACT The sorption of two divalent metals [Pb (II) and Cd (ii)] onto plantain peal waste via kinetic approach has been investigated. The sorption capacity of Cd (II) increases from 0.061 0.189mg/L while Pb (II) increases from 0.071 0.281mg/L, increase in the mass of biomass from 1g 3g decre3ased the adsorption of the metal ions. This may be as a result that high masses of adsorbent donet allow effective contact between the adsorbent and the metal ions. The rate of adsorption increased with decrease in particle size. Pb II and Cd II removal from this study was very rapid within 5 20 minutes to over 50 70% of each metal ion. While examining the bio sorption efficiency, Langmuir and Freundlich models were used. From the Langmuir isotherms, qm which is the measure of maximum adsorption capacity were obtained as 0.050 and 0.198 for Pb II and Cd II, respectively. The adsorption coefficient Kl were obtained as 0.058 and 0.126 for Pb II and Cd II respectively. The separation parameter Sf was less than unity for both metals indicating favourable isotherm. The freundlinch isotherm estimated the adsorption intensity of the sorbate on the sorbent surface. The adsorption intensity 1 /n was obtained as 1.3 and 2.0 for Pb II and Cd II respectively. The Kf value of Pb II was greater than Cd II suggesting that Pb II has greater adsorption intensity towards the biomass than Cd II. However, Pseudo first order model was not adequate to describe the sorption process. Keywords: Sorption conditions, Bio-sorption efficiency models and kinetics. 1. INTRODUCTION Heavy metals are present in the environment [1]. However, various activities by man in recent times have increased the quantity and distribution of heavy metals in the atmosphere, land and water bodies [2]. The extent of this wide spread of heavy metal has become a major threat to plant, animal and human life due to their bioaccumulation tendency and toxicity[3]. Therefore, heavy metal should be removed from municipal and industrial waste waters before discharged into the ambient environment [4]. In pursuit to this however, there technologies for controlling the concentration of these metals in aqueous streams. The conventional technologies which have been used, ranged from granular activated carbon to reverse osmosis [5]. However, these processes are not economically feasible for small scale industries common in developing economies due to huge capital investment [6]. The disadvantages of these conventional methods like incomplete metal removal, high reagent and energy requirements, generation of toxic sludge and so on, has made it imperative to search for alternative adsorbents, which are low cost, simple and sludge free, and environmentally friendly[7]. This present study therefore is aimed at assessing the potentional use of plantain peel waste as an bioadsorbent for the sorption of toxic metals like Pb II and Cd II ions in aqueous media via kinetic approach. 2. MATERIALS AND METHODS Sample Collection A bunch of unripe plantain was collected from Eke Awka market, Awka South Local Government Area, Anambra State. The plantains were washed with deionzed water and air dried. The dried plantain was carefully peeled with a kitchen knife to obtain the plantain peel wastes. The peelings were sun-dried for 8 days. The dried sample was ground using a mechanical grinding and sieved using a manual sieve (standard test sieve ASTME II Specification) to obtain particle sizes of 75um, 150um and 425um. These particle seizes were stored differently in a polyethylene bag for analysis. Activation of Biomass It is often necessary to activate a solid before using it as an adsorbent for sorption studies. The purpose of activation is to increase the surface area of the solid by introducing a suitable degree of porosity into the solid matrix [8]. Again, activation may also produce structural defect on the solid, which may be favourable to sorption processes. The waste plantain peel waste biomass used in the work was chemically activated using hydrochloric acid. The activation process was carried out by mixing 40cm 3 of 1m Hcl with 500g of plantain peel waste in an evaporating dish. The sample was allowed to dry at room temperature. This was done to various particle sizes to be used. 626

Various masses of 1g, 2g and 3g for each of the three particles sizes (75, 150, 425µm) were weighed and kept in a polyethylene away from moisture. Procedure of Adsorption of the Metal Ion Form Aqueous Solution Effect of Metal Ion Concentration Standard solutions of concentration 10, 20, 30 and 40mg/l were made from spectroscopic grade standard of Cd (II) from Cd (NO 3 ) 2 4H 2 O and Pb II from Pb (NO 3 ) 2. 50ml of each metal ion solution was added to accurately weighed (250 ± 1mg) activated biomass in different flasks and agitated for 30mins to ensure that equilibrium was achieved. At the end of the time, the suspension was filtered through whatman No 45 filter paper. The filtered solution was analysed for metal ion by flame atomic absorption spectroscopy (FAAS) model 200A(34) [10]. Effect of Varying Parties Sizes The particle sizes of 75um, l50um and 425um of the activated plantain peel biomass were weighed out 1g, 2g, and 3g in flask l0mls of 10mg/l of standard solution of Cd (NO 3 4H 2 O) was poured into the flask differently and a contact time of 30mins was allowed for adsorption to take place. After the time the suspension was filtered through whatman No 45 filter paper. The procedure was repeated for Pb(NO 3 ) 2 standard solution of (10mg/l). The filtered solution was analysed for metal ion by flame atomic absorption spectroscopy (FAAS) model 200A) [10]. Effect of Contact Time Activated biomass (250 ± 0.01mg) were weighed into several flasks Cd II and Pb II were added to the biomass. The flasks were then labeled for time intervals of 5, 10, 15 and 20mins. The flasks were tightly covered with cellophane and shaken at appropriate time interval, the suspension were filtered using whatman No 45 filter paper. The metal content was determined using FAAS model 200A [10, 11]. Analysis of Metal Content The Cd II and Pb II contents in all experiments were determined with a buck scientific flame Atomic Absorption Spectrophotometer (FAAS) model 200A. Spectroscopic grade standard solution was used to calibrate the instrument. The following wavelengths were used for the metal studied Pb 283.3nm and Cd 228.8nm. Data Evaluation Calculation of the Degree of Metal Ion Removal The amount of Cd II and Pb II ion removed by the biomass during the series of batch investigations were determined using a mass balance equation expressed as in eqn 1 below qe = v/m (co ce) --------------------------------------- (1) Where, qe = Ce = Co = V = M = metal ion concentration on the biomass mg/g biomass an equilibrium. metal ion concentration in solution (mg/l) at equilibrium initial metal ion concentration in solution (mg/l) volume of initial metal ion solution used (l) mass of biomass used (g) Two adsorption models were used to fit the experimental data, the Langmuir and freundilich model. The langmuir (L) equation was chosen for the estimation of maximum adsorption capacity corresponding to complete monolayer coverage on the biomass surface and expressed by eqn 2 q = q m kl c e --------------------------------------------------------- (2) I + kl c e Where kl = langmuir isotherm constant (Lg- 1 ) q m = langmuir monolayer adsorption capacity (mgg 1) The linearized form of the above equation after arrangement is given in eqn 3. c e = 1 + c e ------------------------------------------ (3) qm qmkl q m 627

The experimental data were fitted into equation 3 by plotting c e /q e against c e. Freundilich (f) model was chosen to estimate the adsorption intensity of the sorbent towards the biomass and is represented in eqn 4 Qe = kf(c e )1/n --------------------------------------------------------------- (4) Where qe = the adsorption density (mg of metal ion adsorbed 1g biomass), c e = the concentration of metal ion in solution at equilibrium mg/l Kf and n are freundlich constants. The value of n indicates that affinity of the sorbent towards the biomass. Equation is conveniently used in linear form by taking the natural logarithm of both sides as. Lnq e = in kf + 1/n inc e ---------------------------------------------------- (5) A plot of 1nc e against lnq e that yields a straight line indicated the confirmation of the freundlich adsorption isotherm. The constants 1/n and in kf can be determined from the slope and intercept respectively [11, 12]. Kinetic Treatment of Experimental Data In order to investigate the mechanism of adsorption some equations were applied to the experimental data. The mechanism employed is the pseudo first order mechanism. The kinetics of sorption by biological materials which have been described previously the pseudo first order expression given by langergreen [1] was adopted. The linear form of langergreen pseudo first order model is given by the equation below. In (q e g t ) = in q e k t ------------------------------------------------ (6) Where qe = mass of metal adsorbed at equilibrium (mgg 1) q e = mass of metal adsorbed at tlmgg 1) k = equilibrium rate constant A linear plot of in (q e q t ) versus t conforms the model. However, the actual percentage removal of the metal ions from solution was found to decrease with increase in initial concentration (fig. 1a and 1b). this may be due to the fact that at lower concentration all the ions were adsorbed very quickly and further increases in the initial metal ion concentration leads to the saturation of the surface of biomass. 3. RESULTS AND DISCUSSION 1. Effect of Metal Ion Concentration The experimental result of the uptake of Cd (II) and Pb (II) ions onto the plantain peel waste biomass are at various initial metal ion concentration as shown in fig. 1a & 1b. The sorption capacity of the two metal ions are as follows: The cadmium increases from 0.061 0.189mg/g, that of lead increases from 0.071 0.281mg/g with an increase in concentration of metal ion from 10 40mg/l and a biomass weight of 5g/l. This shows that the adsorbed Pb II is greater than that of Cd II (Pb II > Cd II). Fig. 1a: % METAL ION REMOVED Effect of Concentration on Sorption of Lead (Pb) 628

Fig. 1b: % Metal Ions Removed Effect of Concentration on Sorption of Cadmium (Cd) 2. Effect of Variable Masses and Particle Sizes The experimental result of the uptake of Cd (II) and Pb (II) ions onto the plantain peel waste biomass shows that increase in mass of the biomass from 1g 3g decreases the adsorption of the metal ion. This may be due to the high mass of adsorbent not allowing effective contact between the adsorbent and the metal ions. In the course of the experiment the sorption decreases from 0.381mg/g 0.110mg/g for cadmium and for lead 0.467mg1g 0.146mg/g for particles sizes of 425um as shown in table 2(a). This is applicable to both Cd (II) and Pb (II) ion. Also it shows that Cd (II) ion is much more adsorbed than Pb (II) in all the particle sizes. Comparing the Effect of Particle Sizes on the Rate of Adsorption Human The rate of adsorption increases with decrease in particle size. This is true because the surface area so the adsorbent is increased with smaller particle size, since adsorption is surface phenomenon the rare of adsorption will therefore increase with increased surface area. This is the same for the two metals. Table 1a: Amount of Metal Adsorbed (mg/g) Metal Cd Pb Particle size (um) 425 150 75 425 150 75 1g 0.381 0.426 0.435 0.467 0.467 0.473 2g 0.179 0.199 0.186 0.227 0.231 0.230 3g 0.110 0.214 0.128 0.146 0.148 0.153 Volume 50ml time 30mins conc. 10mg/l Table 1b: Percentage Adsorption of Metal Ions on particle Sizes Metal Cd Pb Particle size masses 425 150 75 425 150 75 1g 79.6 89.1 91.0 97.6 98.1 98.9 2g 75.1 82.5 88.3 95.0 96.4 98.8 3g 69.0 77.6 80.0 90.3 91.8 94.7 Effect of Contact Time Time dependency was conducted in order to obtain how long the plantain peel waste biomass would take to adsorb the metal ions. The data from the time dependent experiment for the removal of the two metal ions by the biomass of the plantain peel waste are presented in Fig. 2a & 2b. As the contact time was increasing from 5 20minutes the amount of metal ions removed by the biomass increased. These data indicate that metal ion removal by the biomass is very rapid for the two metal ions within 5 20 minutes the biomass was capable of removing over 50 70% of each metal ion. It was observed that Pb II ion within the period of 5 20 minutes was much adsorbed than the cadmium II ion. 629

Fig. 2a: Time(mins) Effect of Contact Time on the Sorption of Cadmium (Cd) Time(mins) Fig. 2b: Effect of Contact Time on The Sorption of Lead (Pb) Evaluation of Bio-Sorption Efficiency Sequestering of metallic specie by biomass has been traced mainly into the cell wall of the biomass. The cell wall is not necessarily the only site where the sequestered metal might be situated. They may also be found within the cell, coupled with various organic parts or may crystallize in the cytoplasm [12]. The drying and grinding of bio adsorbent unveil sites where metal ion could be sequestered, increasing the probability of encountering metal ion at such sites. The biosorption data for the removal of Pb II and Cd II were evaluated with langmuir and freuncilich model. 1. Langmuir Isotherm The langmuir isotherm model was chosen for the estimation of maximum adsorption capacity corresponding to complete monolayer coverage on the biomass surface. The plots of specific sorption Ce/qe against the equilibrium concentration Ce for Cd II and Pb II are shown in fig. 3a and 3b, the linear parameters q m and kl are presented in the table 2a below. Table 2: Summary Langmuir Isotherm Cd Pb q m 0.198 0.550 Kl 0.126 0.058 630

The sorption q m which is a measure of maximum adsorption capacity corresponding to complete monolayer coverage showed that plantain peel waste has a high mass capacity for Pb II than Cd II which had q m value of 0.550 and 0.198 respectively. The, adsorption coefficient kl which is related to the apparent energy of sorption of Cd II 0.126 was greater than that of Pb II 0.0587. Further the favourability of adsorption of the two metal ion on the plantain peel waste biomass using the essential feature of the langmuir isotherm model expressed in terms of dimensionless constant called separation factor (sf) [11]. The separation factor is defined by the following relationship. SF = 1 1 + ki Co Where kl = langmuir isotherm constant, Co = initial ion concentration of 9.56 mg/i and 9.66 mg/i for Cd(II) ion and Pb (II) ion respectively. The Sf value of Cd is 0.450 and that of Pb is 0.638 were obtained. The parameters indicate the shape of the isotherm as follows: Sf > 1 unfavourable isotherm Sf 1 linear isotherm Sf 0 irreversible isotherm 0 < Sf < 1 favourable isotherm [11]. The separation parameters for the two metals are less than unity indicating that plantain peel waste biomass is a very good adsorbent for the two metal ions. The Sf value of Pb II ion is greater than that of Cd II ion. Indicating that in a mixed ion system Pb(II) ion will compete for binding site faster than Cd II ion. This observed separation factor indicates that high concentration of Cd II and Pb II ions in an effluent will not be a limiting factor in the ability of plantain waste to absorb metal ions. Fig. 3a: Langmuir Equilibrium Isotherm Model for the Sorption of Cadmium (Cd) On Plantain Peel Waste. 631

Fig. 3b: Ce (mg/l) Langmuir Equilibrium Isotherm Model for the Sorption of Lead (Pb) on Plantain Peel Waste. 2. Freundlich Isotherm The freundlich model was chosen to estimate the adsorption intensity of the sorbate on the sorbent surface. The linear freundlilich isotherm for the sorption of the two divalent metal onto plantain peel waste biomass are presented in fig 4a and 4b. Examination of the plot reveals that freundlich isotherm is also an appropriate model for sorption study of Cd II and Pb II ion. Table 3 shows the linear freundlich sorption isotherm constant. Table 3: Summary Freundlich Isotherm Metal ion Cd Pb Cd II 2.0 0.050 Pb II 1.3 0.038 The kf value of Pb II which is 0.038 is greater than that of Cd II 0.030 suggesting that Pb II had a greater adsorption tendency towards the plantain peel waste biomass than the Cd II. The Freundlich equation parameter. 1/n which is a measure of the adsorption intensity for Cd II is higher than Pb II. Indicating a preferential sorption of Cd II by plantain peel waste biomass. Ince Fig. 4a: Freundlich Equilibrium Isotherm Model for the Sorption of Cadmium (Cd) Plantain Peel Waste. 632

Fig. 4b: Freudilich Equilibrium Isotherm Model for the Sorption of Lead (Pb) on Plantain Peel Waste. Kinetic of Sorption The kinetics of sorption is probably the most important factor in predicting the rate at which sorption takes place for a given system and also very essential in understanding sorber design with sorbate residence time and reactor dimension [11]. However, sorption kinetics shows a large dependence on the physical and/or chemical characteristics of the sorbent material, which also influences the sorption process and the mechanism [12, 13]. Pseudo First Order Model A plot of in (q e q t ) against t gave the pseudo first order kinetics from the plot in fig 5a and 5b, it is observed that the relationship between metal ion diffusivity, in (q e q t ) and time is non linear, indicating that the diffusivity of metal ions onto plantain peel waste biomass surface as film diffusion controlled. The non linearity of the diffusivity plot showed that the pseudo first order equation proposed was not adequate in describing the reaction of the two divalent metal ions on the plantain peel waste biomass surface. It was found that the langergreen equation did not provide a good description for the sorption of the two divalent metal ions. Fig. 5a: Pseudo First Order Plot for Cadmium (Cd). 633

Fig. 5b: Pseudo First Order Plot for Lead (Pb) 4. CONCLUSION The effect of metal ion concentration on adsorption capacities show that plantain (musa x paradisiaca sappientum) peel waste biomass adsorbed metal ions from solution, with an increase in sorption capacity of the biomass with increase metal ion concentration. The actual percent removal of the metal ions from solution decrease with increase in initial metal ion concentration. However, a close look at the data obtained shows that lead is adsorbed more than cadmium using plantain peel waste biomass. Variation in the mass of the adsorbent did not really affect the adsorptivity as such any suitable mass within the range of that used in this research work can be used practically. In addition, the adsorption mechanism for these metal is a stable rapid process and occurred in less than 25 minutes, which implies that adsorption is taking place on the cell wall surface of the plantain peel waste biomass. The equilibrium data fitted the langmuir and freundilich isotherm very well. The separation factor or equilibrium parameter obtained from langmuir isotherm showed that adsorption of metal ions onto the plantain peel waste biomass is favourable. On the whole, the data showed that, plantain peel waste biomass was successful as biosorbent for treating heavy metal contaminated water and may serve as an alternative to conventional means. Hence, not only is musa x paradisiaca sappientum inexpensive and readily available, it also has the potential for metal removal and recovery of metal ions from contaminated water. 5. REFERENCES [1]. Andres M, Y. J. H and Hubert C. J. (1992): Bacterial Biosorption and Retention of Thorium and uranyl cations by myco bacterium smegmatis Journal of radio analyses nuclear letter. Vol. 166. pp 431 440. [2]. Fourest E. and Roux C. J. (1992) Heavy metal biosorption by fungal mycilia by-product. Mechanism and influence of PH. Applied microbiology and biotechnology vol. 37 pp 399 403. [3]. Fris, N and Myers Keith P. (1986) Biosorption of uranium and lead by streptomyces long wood in Botechnology. Bioengineering vol. 28 pp 21 28. [4]. Gadd, G. M and Rome L.D. (1998) Biosorption of copper by fungal melanin. Applied microbiology Biotechnology vol. 29 pp 610 617. [5]. Gang S. and Weixing S. (1998) sunflower as adsorbent for removal of metal ions from waste water. Industrial engineering and chemistry research vol. 37 pp 1324 1328. [6]. Horstall, M. Jnr and Spiff A. I (2004): Kinetic study of divalent metal ion sorption on cadmium biocolor (wild cocoyam) biomass surface Journal of corrosion science and Technology Vol. 2 pp 12 18. [7]. http://www.jbc.org/cgi/content/full/279/25/26028. [8]. Hussein H, Ibrahim S. F, Kandeel, K and Moawad, H. (2004): Biosorption of heavy metals from waste water using pseudomonas specie. Electronic Journal of Biotechnology. Vol. 7 pp 1 11. [9]. Kapoor, A. and Viraragh van, T (1995): Fungal biosorption: an alternative treatment option for heavy metal bearing waste water: A Review Journal of Bioresource. Technology. pp. 6 9. [10]. Kratochril, D and Volesky B. (1998): advances in Biosorption of heavy metals. TIBTESCH vol. 16 pp 291 300. 634

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